Nitrous Oxide Emission from Organic Fertilizer and Controlled Release Fertilizer in Tea Fields

Abstract

A field experiment was conducted for two years in the Green Tea Laboratory of Saitama Prefectural Agriculture and Forestry Research Center, Iruma, Saitama, Japan from March 2014 to December 2015. Controlled release fertilizers (CRF) or organic fertilizers (ORG), which are a mixture of chicken manure and oil cake, were applied with the amount of 450 kg·N·ha⁻¹·year⁻¹ in 2014 and 397 kg·N·ha⁻¹·year⁻¹ in 2015. Nitrous oxide (N₂O) emissions from soil in green tea fields were measured by the closed chamber method. The results showed that CRF has significantly lower N₂O compared to ORG. The cumulative N₂O emissions from CRF accounted for 51% of N₂O emissions from ORG fields and 138% of control with no fertilizer treatment. The N₂O flux from the row was higher than that under the canopy, since fertilizer was applied on the row. However, the total emission from the area between the rows was lower than that under the canopy because the area ratio between the row and canopy was 1:5.

1. Introduction

Tea (Camellia sinensis) is widely cultivated in Japan [1]. To obtain good tea leaf yield and good quality tea, tea fields generally accept a large amount of nitrogen (N) fertilizer in Japan [2] and the N application rate has reached a range of 450–1000 kg·N·ha⁻¹·year⁻¹ [3,4,5]. The high amount of N application rate has led to a large N loss with nitrate (NO₃⁻) leaching, as well as nitrogen dioxide (N₂O) emission [6,7]. Akiyama et al. [8] have reported that the N₂O emission from tea fields in Japan was up to 2.82% ± 1.80% of input N, which is four times higher than that of upland fields, at 0.62% ± 0.48% of input N and nine times greater than paddy fields, at 0.31% ± 0.31%. According to NIES 2012 [9] reports, the N₂O emission from tea fields accounts for approximately 16% of the total N₂O emission from Japanese agricultural fields. Therefore, mitigation of N₂O emission from tea fields in Japan is urgently needed.

To reduce N₂O emission and improve crop N, efficient, controlled-release fertilizer (CRF) has been introduced into many crops [10]. The CRF is coated with polymers, sulfur, or a combination of both [11]. Compared to common chemical fertilizers, which immediately release N into the soil, controlled-release fertilizers and organic fertilizers show various N release patterns and has different N₂O patterns [12]. Quite a number of studies indicate that CRF can mitigate N₂O emission from upland and paddy soils [13,14,15]. However, there is the little information on N₂O emission from tea fields under CRF. Compared to common chemical fertilizer, organic fertilizer (ORG) has a slow N release pattern. Hence, ORG can probably mitigate the N₂O gases emissions due to avoiding high emission peaks [16,17]. Many studies have been conducted to compare N₂O emissions from CRF and common chemical fertilizers in various crop systems [18,19], emphasizing the advantage of CRF to common chemical fertilizers based on the slow release pattern. However, little work has been done to compare N₂O emissions from CRF and ORG.

The tea plant in Japan is cultivated as continuous canopies in rows. The distance between rows of tea plants commonly ranges between 1.5 and 2.0 m. The tea canopy covers a width of 1.0–1.5 m and leaves bare soil between the rows. All fertilizers are applied to the bare soil between the rows of tea plants [20]. No fertilizer is applied to the soil area under the canopy. While the soil in the rows is compacted due to management practices, the soil under the canopy is undisturbed. Higher N₂O flux from the soil under the canopy occurs when there is heavy rainfall [20,21]. The use of CRF is supposed to reduce the N₂O flux for the row, as well as for under the canopy; however, no research has been conducted yet.

Therefore, the aims of this research were: (1) to evaluate the effect of CRF and ORG on N₂O emissions from tea fields; and (2) to evaluate differences in N₂O emissions from soils in rows and under the canopy under different fertilizer applications.

2. Materials and Methods

2.1. Site Description

The study site was located at the Green Tea Laboratory of Saitama Prefectural Agriculture and Forestry Research Center, Iruma, Saitama, Japan (35°80′ N, 139°34′ E). The annual mean air temperature is 14.3 °C, and the total annual precipitation averages 1481.6 mm, considering a 30 year period of observations (1981–2010) by the Japan Meteorological Agency. Tea plant variety Yabukita was planted in 1971. Tea plants were trimmed (spring trimming) on 4 April 2014 and 30 March 2015, and all trimmed leaves and branches were removed from the row, while the leaves and branches that fell into tea bushes remained inside. The tea leaf harvesting times were on 29 May and 15 July in 2014, and on 15 May and 13 July in 2015. The soil was a Silandic Andosol [21]. The basic soil characteristics are shown in

Table 1. Physicochemical characteristics of tea soils.

Location	pH	NH4+-N (mg·kg−1)	NO3−-N (mg·kg−1)	Total C (g·kg−1)	Total N (g·kg−1)	Bulk Density (g·cm−3)
Row	3.63	1.24	6.20	117.6	11.0	0.46
Canopy	3.81	1.74	7.92	104.7	10.5	0.41

Note: NH₄⁺-N and NO₃⁻-N denotes ammonium-nitrogen and nitrate-nitrogen respectively. N, C represent nitrogen and carbon.

.

2.2. Experimental Design

The area of the study site was 832 m² (47 m × 17.7 m) including a buffer 415.8 m². The remaining area was laid out in a randomized complete block design into three treatments with six replications. The length and wide of tea canopy is 11 m and 1.5 m for each plot. The row space was 0.3 m. Both rows along the canopy were fertilized, there were buffer canopies among the treatments. The treatments consisted of no fertilizer as control (denoted as CONT), controlled-released chemical fertilizer (CRF), and organic fertilizer (ORG) treatments. The controlled-released fertilizer in this experiment was sulfur-coated urea (Meister 180-days type, Jcamagri Co., Ltd., Tokyo, Japan), phosphorus (P₂O₅) (Nitto FC Co., Ltd., Nagoya, Japan) and sulfur-coated potash (K₂O) (Meister SOP, Jcam Agri. Co., Ltd., Tokyo, Japan). Organic fertilizers were oil cake (Daiwa Co., Ltd., Hyogo, Japan), and fermented chicken manure (Corporation Omiya Green Service, Omiya, Japan). The nutrition content of organic fertilizer has shown in

Table 2. Chemical component of organic fertilizers.

	N (%)	P (%)	K (%)	C (%)	C/N	Water Content (%)	NH4+-N (mg·kg−1)	NO3−-N (mg·kg−1)	pH
Chickenmanure 2014 & 2015	2.64	5.96	3.95	27.9	10.6	22.4	4.02	0.04	8.1
Oil cake in 2014	12.2	2.56	2.87	20.8	1.70	14.6	16.1	0.83	7.4
Oil cake in 2015	12.1	3.02	3.93	21.6	1.78	14.7	16.0	0.91	7.2

Note: N, P, K, C denotes nitrogen, P₂O₅, K₂O and carbon. C/N means the ratio of carbon and nitrogen, NH₄⁺-N and NO₃⁻-N represents ammonium-nitrogen and nitrate-nitrogen respectively.

. The application rates of N, P₂O₅, and K₂O in each treatment were 450 kg·N·ha⁻¹·year⁻¹, 225 kg·P₂O₅·ha⁻¹·year⁻¹, and 225 kg·K₂O·ha⁻¹·year⁻¹ in 2014, and 397 kg·N·ha⁻¹·year⁻¹, 466 kg·P₂O₅·ha⁻¹·year⁻¹, and 419 kg·K₂O·ha⁻¹·year⁻¹ in 2015. The total amount of fertilizer was split in spring and autumn applications with a rate of 2:1. Fertilizers were applied on 18 March and 2 September in 2014, and on 10 March and 15 September in 2015. All fertilizers were applied as a band application between canopies by incorporation to a depth of 15 cm in soil using a walk-behind rotary tiller.

2.3. Gas Sample Collection and Analysis

The gas sample was conducted by the chamber method. The chambers used in this study comprised a polyvinyl non-transparent circle cylinder with a diameter and height of 20 cm [21]. The bases of the chambers were inserted into the soil between the rows and under the canopies of the tea plants to a depth of 5cm. The bases that had been inserted into the soil between the rows were removed prior to harvesting and fertilizer application, and then returned after the completion of these activities. Vials (20 mL) were vacuumed for 15 min before gas sampling. The 40 mL of air inside the chambers was collected with a 50-mL syringe with a three-way cock. The gas samples in each chamber were collected two times at 20 min intervals, i.e., immediately after the closure of the chamber, and 20 min after placement. Air temperature was measured using an OPTEX thermometer (Optex Co. Ltd., Shiga, Japan) in each chamber.Gas and soil samples were collected once before fertilization and intensively after fertilization. Between fertilizations, gas samples were collected weekly in the growing season and monthly in the winter. The gas samples were taken between 11:00 am and 3:00 pm to measure the daily average gas emission in the field. The N₂O concentration in the air samples were analyzed using a gas chromatograph (GC-2014, Shimadzu, Kyoto, Japan) equipped with an electron capture detector (ECD) held constant at 350 °C. A carrier gas of 5% methane in argon was supplied at a flow rate of 10 mL·min⁻¹. The injection temperature was 80 °C. The gas sampling started from 11 March 2014 to 22 December 2015.

Gas emissions were calculated from the change in the gas concentration in the chamber versus the closure time:

F = ρ × h × (△C/△t) × [273/(273 + T)]

(1)

where F is the gas flux (μg·N·m⁻²·h⁻¹ for N₂O), ρ is the gas density (N₂O-N =1.26 × 10⁹ μm⁻³), h is the height of the chamber from the soil surface (m), △C/△t is the slope of the change of the gas concentration inside the chamber during the sampling period (m³·m⁻³·h⁻¹), and T is the average air temperature during the sampling period (°C).

The emission factor (EF) is defined as the cumulative amount of N₂O emitted from the fertilized treatment minus that from the control treatment and is expressed as a percentage of the N applied [8].

The equation used for the calculation cumulative amount of N₂O is as follows:

$$\mathrm{Cumulative} {\mathrm{N}}_2\mathrm{O} \mathrm{emission}={\sum }_{i=0}^n(R_i\times 24\times D_i)$$

(2)

where R_i is the mean gas flux (mg·N·m⁻²·h⁻¹) of two successive sampling dates, D_i is the number of days in the sampling interval and n is the number of sampling periods.

2.4. Soil Sample Collection and Analysis

Soil temperature was measured at a depth of 10 cm near the chamber. The volumetric soil water content was measured at a depth of 10 cm when the gas samples were collected, using a soil sensor (HydroSense CS 620 sensor, CD 620 display, Cambell Scientific, Inc., Logan, UT, USA). The volumetric soil water content was converted into WFPS using the following formula:

WFPS = Vol/(1 − SBD/2.65)

(3)

where WFPS is the water-filled pore space (%); Vol is the volumetric water content (%); SBD is the soil bulk density (g·cm⁻³); and 2.65 is the soil particle density (g·cm⁻³).

Soil samples were collected from the rows in the different treatments at a depth of 0–10 cm at the same time as the gas sampling. Various physicochemical properties of the soil were measured, including pH, total carbon concentration (TC), total nitrogen (TN), as well as the levels of nitrate (NO₃⁻), and ammonium (NH₄⁺) ions. The procedures used for the laboratory analysis were as follows. The pH of 1:2.5 air-dried soil (weight) to deionized water (volume) (i.e., 20 g soil, 50 mL deionized water) was determined using a glass electrode. The concentrations of NO₃⁻-N and NH₄⁺-N were determined by extracting the mineral N in the soils with a 2 mol·L⁻¹ KCl solution (1:10 soil to KCl solution), which was then filtered through Whatman #42 filter paper and analyzed using a colorimetric method. The absorbance of the extracted solution was measured using a dual wavelength spectrometric method and the indophenol blue method, respectively. For NO₃⁻ concentration, no reagent was added to the 5 mL water samples and measurements were made directly at a wavelength of 220 nm and the absorbance of the extracted solution was measured using a UV-VIS spectrophotometer (Shimadzu UV mini 1240, Shimadzu Corporation, Kyoto, Japan). For NH₄⁺-N analysis, 5 mL of the soil extract, 3 mL of buffer solution, and 2 mL of phenol-nitroprusside were mixed, and the absorbance of the mixed solution was measured after 45 min at a wavelength of 635 nm using a UV–VIS spectrophotometer (Shimadzu UV mini 1240, Shimadzu Corporation, Kyoto, Japan). Solution A contains 16 g of NaOH and 20 mL of NaClO, which is prepared to obtain the final volume of 1 liter by adding distilled water. Solution B contains 30 g Na₂HPO₄12H₂O, 30 g C₆H₅Na₃O₇2H₂O, 3 g EDTA2Na, 60 g phenol, and 0.02 g Na₂ Fe(CN)₅NO2H₂O, which is prepared to obtain a final volume 1 L by adding distilled water. Total carbon and TN were measured using a Sumigraph NC-80 Auto Gas Chromatograph GC-4C device after the soil samples were sieved through a 0.5-mm mesh. The carbon:nitrogen ratio (C:N ratio) of the soil was used in subsequent analyses.

2.5. Statistical Data Analysis

Effects of fertilizer types on cumulative N₂O were compared using a one-way analysis of variance, followed by Tukey’s multiple comparisons test. Relationships between the environmental data and N₂O fluxes were tested by correlation analysis by Pearson’s correlation coefficient, respectively. All statistical analyses were performed using SigmaStat 3.5 statistical software (Systat Software Inc., San Jose, CA, USA). The cumulative amount of N₂O emitted from the tea field was calculated usinga ratio of 1:5 for the row and canopy, corresponding to the row and canopy width.

3. Results

3.1. Environmental Factors

Precipitation occurred intensively during June to September in both years, and the annual precipitation was 814 mm in 2014 and 829 mm in 2015 (Figure 1a). During the hot season (June–September), the mean air temperature was 28.0 °C and the mean soil temperature was 22.7 °C. In the other seasons the mean air temperature was 19.6 °C and 11.9 °C. The highest and lowest air temperatures were 40.1 °C on 7 August and 10.4 °C on 10 March, respectively (Figure 1b). Both soil and air temperatures were higher in rows than under the canopy. The mean WFPS was 20.2% in the soil of the rows and 9.8% in the soil under canopies. The WFPS under the canopy was lower than that of the rows. It started to increase from May until August, and was especially higher in the rainy season in 2015. The WFPS of rows was higher than under the canopies, but not significantly different in both 2014 and 2015. Those of rows were 13.5% and 23.6% in 2014 and 2015, respectively, and 11.4% and 6.5% under the canopies in 2014 and 2015, respectively. The WFPS of both rows and canopies in 2014 were lower than in 2015. Soil pH values in the soil under the canopy was higher than that of soil in the rows from the beginning of the experiment until spring fertilization in 2015, and they were not significantly different (Figure 1d).

There is no significant seasonal change in NH₄⁺-N contents in CONT treatment, and no significant difference found between the NH₄⁺-N contents of rows and under the canopy (p > 0.05) (Figure 2a). The NH₄⁺-N contents in the soil of rows increased rapidly in the soil of rows after fertilizer applications in CRF and ORG treatments (Figure 2b,c).The NH₄⁺-N in the soil of rows were significantly higher than that under the canopy in CRF and ORG treatments (p < 0.05).There was no significant seasonal change in NO₃⁻-N content in CONT treatment (Figure 3a), while there were significant seasonal changes in NO₃⁻-N content during the whole experimental period in both CRF and ORG treatments (Figure 3b,c). The NO₃⁻-N contents in the soil in 2014 did not increase in CRF and ORG treatments after spring and autumn fertilization, while gradually increasing from August, and reaching the highest level on 4 September 2015. There was significant differencein NO₃⁻-N contents in CRF treatment (Figure 3b), but no significant difference for ORG treatment (p > 0.05) (Figure 3c).

3.2. Nitrous Oxide Emission

The N₂O emissions in CONT treatment ranged from −167.9 µg·m⁻²·h⁻¹ to 162.5 µg·m⁻²·h⁻¹ (Figure 4a). Several small emission peaks were observed in July and August 2015. There was no significant difference between the N₂O emission in rows and under the canopy for CONT.There was no high N₂O emission in CRF treatments after spring fertilization and N₂O emission started to increase from the end of June (Figure 4b). After autumn fertilization, a high N₂O emission peak with the value of 475.7 µg·m⁻²·h⁻¹ was observed in 2014 in rows. In 2015, the N₂O emissions in CRF treatment showed similar values with that of the CONT treatment. There was a significant difference between the N₂O emission in rows and under the canopy in CRF treatment. A small N₂O peak from the soil in rows occurred on 2 May and higher emission peaks from soil under the canopy were observed on 4 July in ORG treatment (Figure 4c).The highest amount of N₂O in 2014 was emitted from soil in rows on 8 September, and from soil under the canopy on 17 September. The N₂O emission peaks in ORG treatment gradually decreased from September to October. Nitrous oxide emission gradually increased from soil in rows in ORG treatment just after spring fertilization in 2015, then reached its second highest peak on 17 April with a value of 1161.1 µg·m⁻²·h⁻¹, and then reached the highest peak in the whole experimental period on 24 April, with a value of 1158.0 µg·m⁻²·h⁻¹ (Figure 4c). During the intensive sampling period, which was started in June and ended in late September, N₂O emission peaks were lower in ORG treatment compared with that of CRF treatment. In the whole experimental period, N₂O emission in ORG treatment was significantly higher than that in CONT treatment (p < 0.05), and CRF treatment was not significantly different from CONT and ORG treatments (p > 0.05) (Figure 4a–c).

Nitrous oxide emission was variably correlated with environmental data. In rows, N₂O emission showed positive correlation with NO₃⁻-N concentration (p < 0.05) (

Table 3. Correlation analysis between N₂O emission (µg·N·m⁻²·h⁻¹) and environmental data of the soil.

	NH4+-N (mg·kg−1)		NO3−-N (mg·kg−1)		pH		Air Temp. (°C)		Soil Temp. (°C)		WFPS (%)
	R2	P	R2	P	R2	P	R2	P	R2	P	R2	P
Row	0.50	N.S.	0.02	*	0.61	N.S.	0.22	N.S.	0.64	N.S.	0.97	N.S.
Canopy	0.13	N.S.	0.03	*	0.05	*	0.00	***	0.00	***	0.00	**

Note: NH4⁺-N and NO₃⁻-N denotes ammonium-nitrogen and nitrate-nitrogen; WFPS means water filled pore space; ***, **, *, and N.S. stand for significance at 0.1%, 1%, 5%, and non-significant, respectively.

). For the canopy, N₂O emission showed positive correlations with NO₃⁻-N (p < 0.05), pH, air temperature, soil temperature, and soil moisture at different levels (Table 3).

The annual cumulative N₂O emissions in CRF were 10.8 kg·N·ha⁻¹ and 12.8 kg·N·ha⁻¹ in 2014 and 2015, respectively (Figure 5). The cumulative N₂O emission in 2015 was 11.5% higher than that of 2014. The annual cumulative N₂O emissions were 22.4 kg·N·ha⁻¹ and 30.0 kg·N·ha⁻¹ in 2014 and 2015 in ORG treatment, the cumulative N₂O emission in 2015 was 33.9% higher than that of 2014. In both 2014 and 2015, the cumulative N₂O emissions in ORG treatments were significantly higher than that in CONT and CRF treatments (p < 0.05), while there were no significant differences between CONT and CRF treatments (p > 0.05).

In 2014, the cumulative amounts of N₂O from soil under the canopy were significantly higher in ORG treatment than that of CONT and CRF treatments (Figure 5). Cumulative N₂O emission from the soil in rows was significantly lower in CONT than that of the two fertilized treatments. In 2015, the cumulative N₂O emission from soil under the canopy was significantly higher in ORG treatment than that of CONT and CRF treatments, cumulative N₂O emission from soil in rows in CRF was significantly higher than that in CONT treatment and significantly lower than that in ORG treatment.

In the total two year monitoring period, N₂O emissions were 18.7 kg·N·ha⁻¹, 25.8 kg·N·ha⁻¹, and 52.8 kg·N·ha⁻¹ from CONT, CRF, and ORG, respectively. The N₂O emission factors were 0.84% and 4.03% for CRF and ORG.

4. Discussion

4.1. The Effects of Fertilizer on N₂O Emission

There were more seasonal fluctuations of N₂O emission in ORG treatment compared with that in CONT and CRF treatments (Figure 4). The cumulative N₂O emission from CRF was 51.1% lower than that of ORG. The results from this experiment indicated that CRF could mitigate N₂O emission significantly compared with ORG fertilizer in both years (Figure 5). Coated urea is designed to release N gradually in response to moisture. Water passes by diffusion through pores in the sulfur coating and dissolves the urea, which can then diffuse back into the soil through the intact coating [22,23]. Rupturing of the coating may occur, and increased temperature enhances the rate of N release [24]. In this study, mineral N from the CRF and ORG treatments did not differ significantly throughout the sampling time (Figure 2b,c and Figure 3b,c). These results could be masked by water content and pH factors. Water content and pH are the important regulators to stimulate soil N₂O emission [25]. The chicken manure and oil cake from ORG showed very high water content (22.4% and 14.6%) and pH value (8.1 and 7.4, respectively). The WFPS and pH positively correlated with soil N₂O emission (Table 3).

Although the mineral N in CRF treatment was not significantly lower than that of ORG treatment, cumulative N₂O emission was significantly reduced by applying CRF fertilizer in a two year period (Figure 5).The results of this study are consistent with previous studies. Shoji and Kanno [26] conducted a field study and showed that the peak of N₂O emissions after coated fertilizer application were 18% of the peak of N₂O emission after conventional fertilizer application. As a result, the cumulative N₂O emissions after coated fertilizer application for 70 days were 80% less than the cumulative N₂O emissions after conventional fertilizer application. In this study, the highest peak in CRF treatment was only 475 µg·m⁻²·h⁻¹, while the peak in ORG treatment reached 1161 µg·m⁻²·h⁻¹ during two years of observation. Consequently, the cumulated N₂O emission from controlled-release fertilizer was slightly higher than that of no fertilizer plots, and accounted for just 50% of total N₂O emission from organic fertilizer treatments.

4.2. The Effects of Row and Canopy on N₂O Emissions

In most sampling times, the N₂O emissions from the soil on row were higher than that under the canopy throughout the whole experimental period for all treatments (Figure 4). One of the reasons could be explained by the higher soil and air temperature and soil WFPS in rows than under the canopy (Figure 1) since soil temperature and aerobic conditions are the major factors to regulate soil nitrification and denitrification processes [27,28]. Therefore, CONT with no fertilizer also found higher N₂O emission in rows than that of the canopy. In the case of fertilizer treatments, both NH₄⁺-N and NO₃⁻-N concentrations on rows were higher than that under the canopy in CRF and ORG (Figure 2b and Figure 3b).The higher concentrations of NH₄⁺-N and NO₃⁻-N stimulated more N₂O emissions by providing N sources for nitrification and denitrification processes [27,29]. Furthermore, tea root density under the canopy is higher than that in the rows, and the available N under the canopy is taken up by tea trees more than that of the rows [20]. Thus, the N₂O emissions of rows were significantly higher than that under canopies (Figure 4).

The cumulative amount of N₂O emitted from the tea field was calculated using a ratio of 1:5 for row and canopy, corresponding to the row and canopy width. Thus, even though the emission rate was lower for the canopy, the larger area would lead to the high cumulative amount. Many studies have founded that the canopy can contribute a large amount of N₂O emission [20,21]. Our research also found that N₂O emitted from the soil under the canopy was much higher than for rows (Figure 5). However, the N₂O emitted from the soil under the canopy accounted for 71.7% and 75.2% of the whole emission in CRF in 2014 and 2015, respectively, while it accounted for 83.2% and 52.7%, respectively, for ORG treatments. The significant difference in 2015 could be attributed to fertilizer formats. In CRF, the sulfur coating can improve soil moisture content [10,24,30]. As aresult, the higher N₂O emission would be stimulated by the higher water concentration. From the observation in this research, the WFPS of soil under the canopy was increased 88.8% in 2015 compared with 2014 in CRF treatment, while the WFPS of the soil under the canopy was increased only 44.6% in ORG treatment (data did not showed). Consequently, the percentage of cumulative N₂O emission from the soil under the canopy decreased in 2015 from 83.2% to 52.7% in ORG treatment.

Based on these results, it can be concluded that N₂O emission from the canopy could not be ignored, even if there is no fertilizer applied. Thus, monitoring N₂O emission from the soil under the canopy, as well as from soil between the rows, should be undertaken to determine the precise N₂O emissions from tea fields under different fertilizer types.

5. Conclusions

This study showed that even though both ORG and CRF have slower N release compared to common chemical fertilizer, CRF significantly decreased N₂O emission compared to organic fertilizer in tea fields. The main reason for this was not the release pattern, but the higher water content and pH value of ORG compared to CRF. Physiochemical characteristics of N amendments play a crucial role in controlling N₂O emission from agricultural fields. In this study, we found that row area in tea fields had higher N₂O emission than that of the canopy due to the higher soil temperature, lower moisture, and higher soil mineral N content. However, as the area of the canopy and row was considered, N₂O emitted from the soil under the canopy accounted for over 70% of the whole emission in CRF and 52%–83% of ORG treatments in both years. This indicated N₂O emission from the canopy could not be ignored, even when no fertilizer was applied. In quantification of the N₂O emission from agricultural fields, the area must be categorized in its form of use and the emission must be measured for each form.